Abstract

In this study, various laboratory and field tests were performed to develop an effective automated particle-bound ROS sampling-analysis system. The system uses 2′ 7′-dichlorofluorescin (DCFH) fluorescence method as a nonspecific, general indicator of the particle-bound ROS. A sharp-cut cyclone and a particle-into-liquid sampler (PILS) were used to collect PM2.5 atmospheric particles into slurry produced by a DCFH-HRP solution. The laboratory results show that the DCFH and H2O2 standard solutions could be kept at room temperature for at least three and eight days, respectively. The field test in Rochester, NY, shows that the average ROS concentration was nmol of equivalent H2O2 m−3 of air. The ROS concentrations were observed to be greater after foggy conditions. This study demonstrates the first practical automated sampling-analysis system to measure this ambient particle component.

1. Introduction

Substantial efforts are being made to elucidate the mechanisms of adverse human health effects by airborne particulate matter (PM). Fine particles (PM2.5) have been found to be correlated with cardiopulmonary morbidity and mortality [1]. Ultrafine particles (UFPs, nm) have been associated with effects in animals [2, 3] and humans [4, 5]. However, the chemical components of the particles that drive the mechanisms resulting in health effects are not yet well understood. Since oxidative stress is thought to be a critical factor in driving health effects [1], it is essential to identify and link specific oxidative particulate components, such as reactive oxygen species (ROS).

ROS include oxygen-containing compounds with strong oxidative capacity. Molecules like H2O2, organic peroxides, and nitrite peroxides, ions like hypochlorite ion (OCl−) peroxide anion (), and radicals like hydroxyl () and superoxide radicals (), and organic peroxyl () are all grouped as “reactive oxygen species”. ROS can be generated endogenously during the cell metabolism through reaction of the inhaled PM components such as metals (Fe, Cu, and Zn) and polycyclic aromatic hydrocarbon (PAH) [6, 7]. The excess oxidative stress from the ROS leads to lipid peroxidation, DNA damage, and protein oxidation, and has been implicated in the increased incidence of cardiopulmonary disease, asthma, and chronic obstructive pulmonary disease [8–11]. Recently, ROS was found to be present in PM, especially in the UFPs component [12, 13]. These particle-bound ROS are believed to induce effects on human health analogous to that of endogenous ROS.

The major sources of particle-bound ROS in the atmosphere are reaction between volatile organic compounds (VOC) and oxidants such as ozone (O3) or hydroxyl radicals (OH). For example, the oxidation products of biogenic VOC and O3 have low vapor pressure and can easily condense on the surface of existing PM or nucleate to form secondary organic aerosols (SOA). These components also include peroxides and radical species that constitute some of the particle-bound ROS [14, 15]. In principle, photochemical reactions generate the majority of free radical species in the atmosphere during the daytime. Without sunlight, the particle-bound ROS formation mechanism is largely influenced by the NO3 radical [16] and the OH radical, the latter of which was formed from the ozone and alkene reactions [17]. The specific route through which atmospheric particle-bound ROS are formed remains unclear.

Efforts have been made to characterize the ambient particle-bound ROS. The photochemical intensity was a major factor affecting ROS concentrations in smaller particles, especially in UFPs [18]. The concentration of tropospheric hydroxyl radicals can be described by a linear dependence on solar ultraviolet radiation [19]. Hydroperoxides were simultaneously measured in both gas and aerosol phases, and about 40% of particle-bound H2O2 were associated with PM2.5 [20]. Concentration data on atmospheric ROS in the particle phase are limited and reported in the unit of nmol of equivalent H2O2 m−3 of air [12, 13, 18, 21, 22].

In prior studies, filters were commonly used to manually collect particle-bound ROS. ROS was then extracted from the filters and analyzed using the -dichlorofluorescin (DCFH) fluorescence technique in the laboratory. This method might underestimate ROS concentrations because the short lived species may be more chemically active than the components measured days or weeks later. The method is quite labor intensive [23]. The lack of suitable methods to routinely sample and immediately analyze ROS in the field has restricted the evaluation of the health effects of particle-bound ROS.

A continuous, automated particle-bound ROS system was previously developed [23]. DCFH was employed as a general, nonspecific indicator of particle-bound ROS concentration. A sharp cut cyclone and a particle-into-liquid-sampler (PILS) were used to collect PM2.5 into aqueous slurry that contained the DCFH solution. The fluorescent intensity (FI) was then measured with a flow-through fluorescence detector. Quantification was obtained by relating the sample’s FI to that of an equivalent concentration of H2O2. This initial laboratory system was not deployed because of uncertainties in its operation in the field. Issues of concern included the stability of the reagent solutions under field conditions and the complexity of the design. The current study presents the results from the laboratory testing of a modified system and measurement of the solution stabilities leading to field measurements of atmospheric particle-bound ROS concentrations in Rochester, NY.

2. Experimental

2.1. Instruments

A schematic diagram of the automated sampling-analysis system is shown in Figure 1. The detailed design and construction of the system were introduced in the previous study [23]. During the optimization and laboratory testing of the system, the membrane reactor and superserpentine reactor were found not to significantly improve the reaction among the DCFH, horseradish peroxidase (HRP) and ROS. Therefore, they were removed from the system and the HRP was directly dissolved into the DCFH solution.

The current system included a PM2.5 sharp-cut cyclone, a manganese dioxide (MnO2) denuder to remove gas phase oxidants, and a particle-into-liquid-sampler (PILS, Metrohm Inc.) as the inlet system. The solutions are circulated using an 8-channel peristaltic pump through a selection valve, and a fluorescence detector (FP2020, Jasco Inc.). The sample and blank cycles were run for 3 minutes and 7 minutes, respectively, via the selection valve to eliminate effects of one cycle on the next. To minimize variability arising by visible and long-wavelength UV radiation, as well as to prevent photo-oxidation of the DCFH, the flow lines were covered with aluminum foil. The sampling flow rate was 16.7 L/min.

2.2. Reagents

Two solutions, DCFH with HRP and H2O2 standards, were prepared in a dark environment before the measurements. DCFH is a nonfluorescent reagent that becomes fluorescent upon reaction with ROS. Glass containers were wrapped with aluminum foil to prevent exposure to light. All solutions were prepared with high purity water (resistivity: 18.2 MΩ·cm at 25°C, Millipore Corp.).

The DCFH and HRP solutions were prepared at 5 μM and 0.5 units/mL, respectively, as described in Appendix A. An standard H2O2 solution was used to develop the calibration curve. The specific preparation process of H2O2 standards through a series of dilutions of 30% H2O2 is shown in Figure 2. Final H2O2 concentrations of , , , M were made by mixing 0.1 mL of intermediate H2O2 solutions of M, M, M, and M with 3 mL DCFH solution prepared with HRP. Standard curves were developed from measuring the FI of these final four concentrations of H2O2.

Figure 2: Standard H2O2 preparation process.

2.3. Procedure

The standard operation procedure for running the automated ROS system is given in Appendix B. Calibration of the system was performed with standard H2O2 solutions of concentrations ranging from 100 to 400 nM, prepared by serial dilutions of a 30% stock solution of H2O2, with MilliQ water serving as a blank. A HEPA filter was placed in front of the system during calibration running. Figure 3 shows the blank-subtracted linear calibration curve obtained in the field. The system was linear () over the range of H2O2 concentrations by least-squares analysis. The relationship between H2O2 concentration and FI is expressed as the equation in the figure.

Figure 3: Calibration plot of the system with standard H2O2 solutions in the field.

2.4. Sampling Location

The particle-bound ROS concentrations, O3 concentrations and meteorological parameters (ambient temperature, relative humidity, wind direction and speed) were continuously measured during the period of August 12 to 18, 2009 at the New York State Department of Environmental Conservation (NYSDEC) site in Rochester, NY. The site is located at N, W, adjacent to Interstate Highway I-490 and I-590, as well as NY Route 96, a major route carrying traffic traveling to and from downtown Rochester (see Figure 4).

Figure 4: Location of the sampling site in Rochester, NY.

3. Results and Discussion

3.1. Stabilities of the DCFH and H2O2 Solutions

The stability of the chemical reagents is important for a practical system that can be maintained in the field with a reasonable level of effort. Therefore, the stabilities of DCFH and H2O2 standards were examined. The experimental stability results for 5 μM DCFH stored at room temperature are presented in Figure 5 and Table 1. It can be seen that 5 μM DCFH was stable for three days at room temperature. The stability of the H2O2 standards is shown in Figure 6 and Table 2. The solutions can be kept at room temperature for up to eight days. These results provide the feasibility in the field deployment of the automated sampling-analysis system since the unit does not require daily solution preparation.

3.2. Laboratory Testing of the System

Laboratory tests were performed by sampling particle-bound ROS from an α-pinene-ozone generator [24] for 30 minutes at a flow rate of 16.7 L min−1. The continuous sample and filter sample were compared with H2O2 standard solutions (see Figure 7). During a 30-minute sampling period, the FI was constant. The filter point represents sample taken on a baked quartz filter for 15 minute intervals. This sample duration limits the loss of short lifetime ROS. 50 mL of 5 μM DCFH was added to the filter sample and the filter was then sonicated for another 15 minutes. The FI of the filter particle-bound ROS was comparable to that measured with the continuous system. The FI results of filter and continuous samples were plotted in the standard calibration curve shown in Figure 7.

A somewhat higher FI was obtained from the filter sample, which contradicts the assumption that the filter sampling method may result in the loss of short lifetime ROS, leading to lower FI in filter sample than from continuous system sample [23]. The 15-minute extraction of the filter sample probably increased the extent of DCFH oxidization rather than decreased short lifetime ROS. Another possible reason was that the extraction volume of DCFH solution was 50 mL, which was larger than the volume used for the continuous system sample (10 mL). Therefore, higher FI for filter particle-bound ROS was produced. After the chemical reagents stability check and laboratory performance testing, the automated particle-bound ROS sampling-analysis system was ready for field testing.

3.3. Field Testing of the System

Table 3 summarizes statistics of meteorological parameters. Persistently sunny and humid weather (average ambient temperature: 25.75°C, average relative humidity: 66.17%) was given by Ontario Lake seated to the north. The prevailing winds during this period were mainly from the southwest with an average wind speed of 1.44 m/s. During the seven days of study, there was one foggy day (6:00–9:00 AM on August 13) and two rainy days (precipitation less than 0.4 cm and lasted for only five minutes).

Figure 8 shows the diurnal variations of hourly average particle-bound ROS concentrations measured on both weekdays and weekend days. The weekday concentrations were generally higher than those measured on weekends. The greatest difference was observed during early morning when primary emissions from motor vehicles operating on nearby highways (I-490 and I-590). There were significant differences in traffic volumes between weekdays and weekend days. The highest average ROS concentrations occurred during the afternoon. The daytime ROS concentrations were slightly greater than the nighttime levels on both weekdays and weekends.

Similar results have been found in Rubidoux, CA, and New York City, where the particle-bound ROS did not drop as much as the O3 concentrations during nighttime [12, 13]. New formation through the NO3 pathway and the transported longer-lived ROS play important roles in the elevated nighttime ROS concentrations. The nitrate radical reactions along with the oxidation of alkenes by the residual ozone led to ROS concentrations that were only slightly lower than the daytime concentrations [22]. These diurnal patterns suggest that photochemical reactions and vehicular emissions are the main sources of the atmospheric particle-bound ROS in urban areas.

Table 4 compares the particle-bound ROS concentrations measured in different urban locations with filter collection and extraction methods. Except for the flushing, NY study, all of the studies were conducted during the summer. The overall average ROS concentration from all the studies was 6.1 nmol m−3. The lowest ROS concentration (0.54 nmol m−3) was measured in Taipei, Taiwan, which was an order of magnitude lower than the ROS concentrations in the other studies. Short-lived ROS with lifetime less than 3-hr cannot be estimated, since 3-hr samples were collected in that study [22]. Thus, concentrations of ROS with lifetime less than 3-hr might be greatly underestimated. The average particle-bound ROS concentration of 8.3 ± 2.2 nmol m−3 measured in this study is among the typical values reported for the urban sites of U.S. and Asia.

Table 4: Summary of previous particle-bound ROS studies.

Table 5 summarizes the Pearson correlation coefficients between the hourly averaged ROS values, the other measured pollutants, and the meteorological variables. All the variables were measured at the same site and were averaged to hourly values. Details of the measurements are described elsewhere [25–27]. The scatter plot of the average ozone concentrations and the corresponding ROS concentrations for the entire sampling period is shown in Figure 9. The ozone concentrations, measured as a potential indicator of the intensity of photochemical reactions [18], were obtained from standard photometric ozone monitors maintained by the NYSDEC at this location. The statistically high correlation () between ozone and ROS concentrations indicates that the formation of ROS is strongly influenced by photochemical activity, consistent with the previous studies [13, 18, 22].

The largest standard deviation of ROS concentration was found for the highest level shown as the top point. It was due to the higher ROS concentrations measured on the August 13, a foggy morning, with an average ROS concentration of 12.31 nmol m−3. This event may have resulted from rapid uptake of water-soluble oxidants into the aqueous phase leading to high residual ROS concentration. In addition, the yields of H2O2 and other complex peroxides were observed to increase substantially in the presence of water vapor in the air from another recent study [28].

4. Conclusions

Chemical reagent stability and laboratory performance testing suggested the feasibility of field application of an automated atmospheric particle-bound ROS sampling-analysis system. Sampling of summertime ambient ROS was successfully performed for seven days in Rochester, NY. The average ROS concentration of 8.3 ± 2.2 nmol m−3 is among the typical values reported for the urban sites in the U.S. and Asia. It was also found that photochemical reactions and vehicular emissions were two major factors affecting the particle-bound ROS concentrations in urban atmosphere. Nighttime ROS concentrations were only slightly lower than daytime levels. The ROS concentrations were observed to be greater in and after foggy weather conditions than clear days. It is probably because there was uptake or production of oxidants in the aqueous phase and when the water evaporated, it left significant amounts of residual ROS in the atmosphere.

This study has produced the first practical system to measure this particle component. Uncertainties including the PILS particle capture efficiency, the denuder gas-phase ROS removal efficiency, and the denuder replacement frequency need to be quantified in future experiments. The automated particle-bound ROS sampling-analysis system could conceivably be useful for regulatory communities to control ROS pollution. Further studies are required to use ROS concentrations measured at different locations in different seasons and relate them to human cardiopulmonary diseases.

B. Standard Operating Procedure for the ROS Monitor

The standard operation procedure for running the automated ROS system is the following. (i)Check connections between each unit and all tubing to ensure no leakage.(ii)Turn on the sampling pump and the air dryer and make sure the sampling flow rate at 16.7 L/min.(iii)Turn on the peristaltic pump, and set the rotation rate at 35 rotations per minute. (iv)Turn on the PILS and set the tip temperature at 100°C. (v)The PILS steam generator temperature will reach 150°C with the setting temperature at 100°C. Subsequently, turn on the fluorescence detector, and set the gain at 1000, attenuation at 1, response speed at standard, excitation and emission wavelength at 485 and 530 nm, respectively. (vi)Start the computer, set the sampling period of 3 minutes and rinsing period of 7 minutes. (vii)Start the “Logger Lite” software (version 1.3.2, Vernier Software & Technology) and build a file to save the data.

Acknowledgments

This work was supported by the United States Environmental Protection Agency (EPA) through Science to Achieve Results (STAR) Grant no. RD83107801, a Syracuse Center of Excellence CARTI Project Award, which is supported by a grant from the U.S. Environmental Protection Agency [Award no. X-83232501-0], the Electric Power Research Institute under Agreement no. W06325, and the New York State Energy Research and Development Authority (NYSERDA) through Contracts nos. 8650 and 10604. Although the research described in this paper has been funded wholly or in part by the EPA, it has not been subjected to the Agency's peer and policy review and, therefore, does not necessarily reflect the views of the Agency and no official endorsement should be inferred.